Toxic cyanobacterial breakthrough and accumulation in a drinking water plant: A monitoring and treatment challenge

École Polytechnique de Montreal, Civil, Mineral and Mining Engineering Department, P.O. Box 6079, Station Centre-ville, Montreal, Quebec, Canada.
Water Research (Impact Factor: 5.53). 11/2011; 46(5):1511-23. DOI: 10.1016/j.watres.2011.11.012
Source: PubMed


The detection of cyanobacteria and their associated toxins has intensified in recent years in both drinking water sources and the raw water of drinking water treatment plants (DWTPs). The objectives of this study were to: 1) estimate the breakthrough and accumulation of toxic cyanobacteria in water, scums and sludge inside a DWTP, and 2) to determine whether chlorination can be an efficient barrier to the prevention of cyanotoxin breakthrough in drinking water. In a full scale DWTP, the fate of cyanobacteria and their associated toxins was studied after the addition of coagulant and powdered activated carbon, post clarification, within the clarifier sludge bed, after filtration and final chlorination. Elevated cyanobacterial cell numbers (4.7 × 10(6)cells/mL) and total microcystins concentrations (up to 10 mg/L) accumulated in the clarifiers of the treatment plant. Breakthrough of cells and toxins in filtered water was observed. Also, a total microcystins concentration of 2.47 μg/L was measured in chlorinated drinking water. Cyanobacterial cells and toxins from environmental bloom samples were more resistant to chlorination than results obtained using laboratory cultured cells and dissolved standard toxins.

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    • "SYTO9 marking all cell membranes and propidium iodide (PI) binding only cells with lethally damaged membranes (Boulos et al., 1999; Stocks, 2004; Berney et al., 2007). Cyanotoxin analyses were conducted via an online solid phase extraction-liquid chromatography coupled to tandem mass spectrometry (online SPE-LC-MS/MS) as previously described by Zamyadi et al. (2012b) "
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    ABSTRACT: Intense accumulation of toxic cyanobacteria cells inside plants, unsuccessful removal of cells and consequent breakthrough of cells and toxins into treated water have been increasingly documented. Removal or destabilisation of cells in the pre-treatment stage using pre-ozonation could be an efficient practice as ozonation has been proven to be effective for the removal of cells and toxins. However, several unknowns including the ozone demand, the potential release of cell-bound toxins and organic matter and their impact on treatment train needs to be addressed. The general objective of this work was to study the impact of direct ozonation on different potentially toxic cyanobacteria genera from natural blooms. Water samples from five cyanobacterial bloom events in Lake Champlain (Canada) were ozonated using 2e5 mg/L O 3 for a contact time of maximum 10 min. Cyanobacterial taxonomic enumeration, cyanotoxins, organic matter and post-chlorination disinfection by-product formation potential analyses were conducted on all samples. Anabaena, Aphanizomenon, Microcystis and Pseudanabaena were detected in bloom water samples. Total cell numbers varied between 197,000 and 1,282,000 cells/mL prior to ozonation. Direct ozonation lysed (reduction in total cell numbers) 41%e80% of cells and reduced released toxins to below detection limits. Microcystis was the genus the least affected by ozonation. However, DOC releases of 0.6e3.5 mg/L were observed leading to maximum 86.92 mg/L and 61.56 mg/L additional total THMs (four trihalomethanes) and HAA 6 (six haloacetic acids) formation, respectively. The results of this study demonstrate that vigilant application of pre-ozonation under certain treatment conditions would help to avoid extreme toxic cells accumulation within water treatment plants. ScienceDirect journal homepage: ww w.else /wa tres w a t e r r e s e a r c h 7 3 (2 0 1 5) 2 0 4 e2 1 5
    Water Research 01/2015; 73:204-215. DOI:10.1016/j.watres.2015.01.029 · 5.53 Impact Factor
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    • "Cyanobacteria represent one of the major causes of ecosystem degradation and impairment of the economical value of freshwater resources. Specific strains produce a wide range of powerful toxins, with important implications for health risks associated with the human exploitation of recreational and drinking waters (Meriluoto and Codd, 2005; Mankiewicz-Boczek et al., 2011; Zamyadi et al., 2012). The principal classes of cyanotoxins are microcystins, nodularins, anatoxin-a and homoanatoxin-a, anatoxin-a(S), saxitoxins and cylindrospermopsins (Metcalf and Codd, 2012; M ejean et al., 2014). "
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    ABSTRACT: In order to identify the cyanobacterial species responsible of anatoxin-a (ATX) production in Lake Garda (Northern Italy), an intensive isolation and culturing of filamentous cyanobacteria were established since 2014 from environmental samples. In this work, we report a detailed account of the strategy adopted, which led to the discovery of a new unexpected producer of ATX, Tychonema bourrellyi. So far, this species is the first documented example of cultured Oscillatoriales able to produce ATX isolated from pelagic freshwater ecosystems. The isolated filaments were identified adopting a polyphasic approach, which included microscopic species identification, genetic characterisation and phylogenetic analyses based on 16S rRNA genes. The taxonomic identification was further confirmed by the high (>99%) rbcLX sequence similarities of the T. bourrellyi strains of Lake Garda with those deposited in DNA sequence databases. More than half of the isolates were shown to produce a significant amount of ATX, with cell quota ranging between 0.1 and 2.6 µg mm-3, and 0.01 and 0.35 pg cell-1. The toxic isolates were tested positive for anaC of the anatoxin-a synthetase (ana) gene cluster. These findings were confirmed with the discovery of one ATX producing T. bourrellyi strain isolated in Norway. This strain and a further non-ATX producing Norwegian T. bornetii strain tested positive for the presence of the anaF gene of the ana gene cluster. Conversely, none of the Italian and Norwegian Tychonema strains were positive for microcystins (MCs), which was also confirmed by the absence of mcyE PCR products in all the samples analysed. This work suggests that the only reliable strategy to identify cyanotoxins producers should be based on the isolation of strains and their identification with a polyphasic approach associated to a concurrent metabolomic profiling.
    Water Research 11/2014; 69:68-79. DOI:10.1016/j.watres.2014.11.006 · 5.53 Impact Factor
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    • "MC concentrations vary greatly in different water resources , ranging from microgram per liter to milligram per liter (Zamyadi et al., 2012a, b). To ensure drinking water safety, the World Health Organization (WHO) has recommended a guideline value of 1.0 mg/L for MC-LR in drinking water (WHO, 2004). "
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    ABSTRACT: The intermediates and byproducts formed during the ozonation of microcystin-LR (MC-LR, m/z = 995.5) and the probable degradation pathway were investigated at different initial molar ratios of ozone to MC-LR ([O3]0/[MC-LR]0). Seven reaction intermediates with m/z ≥ 795.4 were observed by LC/MS, and four of them (m/z = 815.4, 827.3, 853.3 and 855.3) have not been previously reported. Meanwhile, six aldehyde-based byproducts with molecular weights of 30-160 were detected for the first time. Intermediates structures demonstrated that ozone reacted with two sites of MC-LR: the diene bonds in the Adda side chain and the Mdha amino acid in the cyclic structure. The fragment from the Adda side chain oxidative cleavage could be further oxidized to an aldehyde with a molecular weight of 160 at low [O3]0/[MC-LR]0. Meanwhile, the polypeptide structure of MC-LR was difficult to be further oxidized, unless [O3]0/[MC-LR]0 > 10. After further oxidation of the intermediates, five other aldehyde-based byproducts were detected by GC/MS: formaldehyde, acetaldehyde, isovaleraldehyde, glyoxal and methylglyoxal. Formaldehyde, isovaleraldehyde and methylglyoxal were the dominant species. The yields of the aldehydes varied greatly, depending on the value of [O3]0/[MC-LR]0.
    Water Research 06/2014; 63C:52-61. DOI:10.1016/j.watres.2014.06.007 · 5.53 Impact Factor
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